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The International Collaboration on Air Pollution and Pregnancy Outcomes: Initial Results

[do action=”authors”]Jennifer D. Parker1, David Q. Rich2, Svetlana V. Glinianaia3, Jong Han Leem4, Daniel Wartenberg5, Michelle L. Bell6, Matteo Bonzini7, Michael Brauer8, Lyndsey Darrow9, Ulrike Gehring10, Nelson Gouveia11, Paolo Grillo12, Eunhee Ha13, Edith H. van den Hooven14,15, Bin Jalaludin16, Bill M. Jesdale17, Johanna Lepeule18,19, Rachel Morello-Frosch17,20, Geoffrey G. Morgan21,22, Rémy Slama18,19, Frank H. Pierik15, Angela Cecilia Pesatori23, Sheela Sathyanarayana24, Juhee Seo13, Matthew Strickland9, Lillian Tamburic25, Tracey J. Woodruff26[/do][do action=”affiliations”]1 National Center for Health Statistics, Centers for Disease Control and Prevention, Hyattsville, Maryland, USA, 2 Department of Community and Preventive Medicine, University of Rochester School of Medicine and Dentistry,Rochester, New York, USA, 3 Institute of Health and Society, Newcastle University, Newcastle upon Tyne, England, United Kingdom, 4 Department of Occupational and Environmental Medicine, Inha University, Incheon, Republic of Korea, 5 UMDNJ-Robert Wood Johnson Medical School, Piscataway, New Jersey, USA, 6 Yale University, School of Forestry and Environmental Studies, New Haven, Connecticut, USA, 7 Department of Experimental Medicine, University of Insubria, Varese, Italy, 8 University of British Columbia, Department of Medicine, Vancouver, British Columbia, Canada, 9 Department of Environmental Health, Emory University, Atlanta, Georgia, USA, 10 Institute for Risk Assessment Sciences, Utrecht University, Utrecht, the Netherlands, 11 Department of Preventive Medicine, School of Medicine of the University of São Paulo, São Paulo, Brasil, 12 Epidemiology Unite, “Fondazione IRCCS Ca’Granda—Ospedale Maggiore Policlinico,” Milan, Italy, 13 Department of Preventive Medicine, Ewha Womans University, Seoul, Republic of Korea, 14 Generation R Study Group, Erasmus Medical Center, Rotterdam, the Netherlands, 15 Department of Urban Environment, Netherlands Organisation for Applied Scientific Research (TNO), Delft, the Netherlands, 16 Centre for Research, Evidence Management and Surveillance, Sydney South West Area Health Service, and School of Public Health and Community Medicine, University of New South Wales, Sydney, Australia, 17 Department of Environmental Science, Policy and Management, University of California–Berkeley, Berkeley, California, USA, 18 INSERM, Team of Environmental Epidemiology applied to Reproduction and Respiratory Health, U823, Institut Albert Bonniot, Grenoble, France., 19 University J. Fourier Grenoble, Grenoble, France, 20 School of Public Health, University of California–Berkeley, Berkeley, California, USA, 21 North Coast Area Health Service, Lismore, New South Wales, Australia, 22 University Centre for Rural Health–North Coast, University of Sydney, Sydney, New South Wales, Australia, 23 Department of Occupational and Environmental Health, Università di Milano, Milan, Italy, 24 Seattle Children’s Research Institute, University of Washington, Seattle, Washington, USA, 25 University of British Columbia, Centre for Health Services and Policy Research, Vancouver, British Columbia, Canada, 26 Center for Reproductive Health and the Environment. University of California–San Francisco, San Francisco, California, USA[/do][do action=”citation-string”]Environ Health Perspect 119:1023-1028 (2011). [online 09 February 2011] [/do]

Research Article


[do action=”abstract”]

Background: The findings of prior studies of air pollution effects on adverse birth outcomes are difficult to synthesize because of differences in study design.

Objectives: The International Collaboration on Air Pollution and Pregnancy Outcomes was formed to understand how differences in research methods contribute to variations in findings. We initiated a feasibility study to a) assess the ability of geographically diverse research groups to analyze their data sets using a common protocol and b) perform location-specific analyses of air pollution effects on birth weight using a standardized statistical approach.

Methods: Fourteen research groups from nine countries participated. We developed a protocol to estimate odds ratios (ORs) for the association between particulate matter ≤ 10 μm in aerodynamic diameter (PM10) and low birth weight (LBW) among term births, adjusted first for socioeconomic status (SES) and second for additional location-specific variables.

Results: Among locations with data for the PM10 analysis, ORs estimating the relative risk of term LBW associated with a 10-μg/m3 increase in average PM10 concentration during pregnancy, adjusted for SES, ranged from 0.63 [95% confidence interval (CI), 0.30–1.35] for the Netherlands to 1.15 (95% CI, 0.61–2.18) for Vancouver, with six research groups reporting statistically significant adverse associations. We found evidence of statistically significant heterogeneity in estimated effects among locations.

Conclusions: Variability in PM10–LBW relationships among study locations remained despite use of a common statistical approach. A more detailed meta-analysis and use of more complex protocols for future analysis may uncover reasons for heterogeneity across locations. However, our findings confirm the potential for a diverse group of researchers to analyze their data in a standardized way to improve understanding of air pollution effects on birth outcomes.

[/do][do action=”abstract”]Key words: air pollution, birth weight, ICAPPO, low birth weight, particulate matter, pregnancy[/do]

[do action=”notes-rule-above”]Address correspondence to J.D. Parker, National Center for Health Statistics, 3311 Toledo Rd., Room 6107, Hyattsville, MD 20782 USA. Telephone: (301) 458-4419. Fax: (301) 458-4038. E-mail:[/do][do action=”notes”]M.L.B. was supported in part by National Institutes of Health grant 1R01ES016317. J.L. was supported by a postdoctoral grant from Institut national de la santé et de la recherche médicale (INSERM). U.G. was supported by a research fellowship of the Netherlands Organization for Scientific Research (NWO).[/do][do action=”notes”]The authors declare they have no actual or potential competing financial interests.[/do][do action=”notes”] Received 15 July 2010; accepted 09 February 2011; online 09 February 2011.[/do]

[do action=”notes”] The findings and conclusions in this article are those of the authors and do not necessarily represent the views of the National Center for Health Statistics, Centers for Disease Control and Prevention. [/do]

Evidence that poor air quality can adversely affect birth outcomes is increasing. A small number of review articles have summarized existing studies and concluded that there is likely an adverse effect of air pollution on pregnancy outcome (Glinianaia et al. 2004; Ritz and Wilhelm 2008; Šrám et al. 2005). However, estimated associations between these outcomes and air pollutant exposures over the whole pregnancy and during specific time windows (e.g., trimester of pregnancy) have been inconsistent, making definitive conclusions difficult (Glinianaia et al. 2004; Slama et al. 2008; Woodruff et al. 2009).

Comparisons of findings across different geographic locations are hindered, in part, by differences in research designs. Although most published studies have reported adverse pregnancy outcomes in association with prenatal exposure to air pollution, inconsistent findings reported by some studies prompted a series of workshops to discuss this relatively new area of investigation (Slama et al. 2008; Woodruff et al. 2009) and the formation of the International Collaboration on Air Pollution and Pregnancy Outcomes (ICAPPO) (Woodruff et al. 2010). The primary objective of ICAPPO is to understand how differences in research design and methods contribute to variations in findings.

As part of this effort, a feasibility study was developed to determine whether it would be possible to use a common protocol to reanalyze existing data sets that were created to answer similar but not identical research questions. A workshop was held in Dublin (25–29 August 2009) to share and discuss the initial results of the feasibility study. In this report, we describe the common research protocol and participating studies. Throughout this article, study results from each research group are referred to by name [e.g., EDEN study (Etude des Déterminants pré et post natals du développement et de la santé de l’Enfant)] if available, otherwise by location (e.g., Seattle study). Additionally, we present estimated odds ratios (ORs) for the association between low birth weight (LBW) among term births and exposure to ambient particulate matter with an aerodynamic diameter ≤ 10 μm (PM10) during pregnancy.


Through discussion with the larger group of ICAPPO participants and detailed planning by a smaller group (J.D.P., D.Q.R., S.V.G., J.H.L.), a protocol for the feasibility study was developed, agreed upon, and distributed to a geographically diverse group of researchers. To maximize the number of participating groups, we deliberately simplified the protocol by restricting the primary statistical analysis to one outcome (LBW in term births) and the air pollution exposure (PM10) available for the largest number locations (Woodruff et al. 2010).

Cohort restrictions. We limited the study to live-born, singleton, term (37–42 complete weeks of gestation) infants with known birth weight, maternal education [or another measure of socioeconomic status (SES)], dates of birth and conception (often based on last menstrual period), and ambient PM concentrations, as described below, during pregnancy. The primary outcome was term LBW, defined as birth weight < 2,500 g.

Air pollution exposure. The primary exposure variable was the ambient concentration of PM10 averaged over the entire pregnancy. PM10 concentrations were assigned to each subject using the approach employed by each research group in their original work. Although we focused on PM10, investigators also were encouraged to provide results for fine PM [≤ 2.5 μm in aerodynamic diameter (PM2.5)] if available. Studies without PM10 data provided effect estimates for PM2.5 or black smoke exposures during pregnancy.

Black smoke approximates PM4 (< 4 µm in diameter) (Muir and Laxen 1995); results for black smoke are presented alongside the PM10 results for the PAMPER (Particulate Matter and Perinatal Events Research) study (Newcastle upon Tyne, UK). The methods for modeling the PAMPER black smoke exposures are described elsewhere (Fanshawe et al. 2008).

Socioeconomic status. ICAPPO participants identified SES as a potentially important control variable when assessing pollution and birth outcomes (Slama et al. 2008; Woodruff et al. 2009) and agreed to use maternal education as the primary measure of SES in the feasibility study. Maternal education is commonly used as an SES measure in perinatal studies and has been shown to be related, albeit imperfectly, with other measures of SES (Kaufman et al. 2008; Parker et al. 1994; Pickett et al. 2002). If maternal education was unavailable, using different individual or area-level SES measures was allowed. Because the collection and meaning of maternal education for these studies differ among the study locations, its form as an analytic covariate differed among the study locations.

Other covariates. Participants also were encouraged to provide estimates adjusted for additional covariates as described below. Although additional variables make comparisons of results across locations more challenging, they allowed us to examine how additional adjustments specific to each location might influence estimates reported by each study.

Primary statistical analysis. We used logistic regression, with term LBW as the dependent variable and PM10 as a continuous explanatory variable; black smoke was used in the PAMPER study, as described above. Results are reported as ORs per 10-μg/m3 increase in average concentration during pregnancy to facilitate synthesis of results. Results from two models were examined: Model 1 covariates were PM10 and study-specific maternal education or other SES measure; model 2 covariates were PM10, maternal education or other SES measure, plus other study location–specific covariates as described above.

Secondary statistical analyses. For these analyses, we suggested modeling continuous term birth weight as an outcome (using linear regression) and/or using PM2.5 as an exposure measure. In addition, results from models describing associations after controlling for different SES measures were contributed. Secondary analyses were encouraged but not required for participation, so results of secondary analyses were not reported by all investigators.

Although full meta-analyses were not performed, in our examination of results, initial tests of homogeneity across study locations were conducted using fixed-effects models (Sterne et al. 2001). In these tests, the null hypothesis of homogeneity was rejected with p-values < 0.05.


Locations. Fourteen research groups from nine countries participated (Table 1). Of these, six reported results for PM10 only, six for both PM10 and PM2.5, one for PM2.5 only (Seattle study), and one for black smoke only (PAMPER study). Most data were from the late 1990s to the mid-2000s. However, the PAMPER study comprised births from 1962 through 1992. The number of eligible births ranged from slightly > 1,000 in the EDEN study, Nancy and Poitiers, France] to > 1 million in the California study, although there was some variability within studies depending on the exposure measure and covariates. The percentage of LBW among term births ranged from 1.15% in the PIAMA (Prevention and Incidence of Asthma and Mite Allergy) study (Netherlands) to 3.77% in the São Paulo study (Table 1).

Table 1: Birth years, number of births, percent term LBW,<br />         and measure of SES used in model 1 (adjusted for SES only), by<br />         study.

Table 1

Birth years, number of births, percent term LBW, and measure of SES used in model 1 (adjusted for SES only), by study.

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By design, data sets used in the feasibility study have been used for previous studies of pollution and pregnancy outcomes or are intended for such use. However, these are not necessarily studies of PM10 or term LBW, and previously published results may have been based on earlier versions of study data sets (Bell et al. 2007, 2008; Brauer et al. 2008; Darrow et al. 2009a, 2009b; Gehring et al. 2011; Glinianaia et al. 2008; Gouveia et al. 2004; Ha et al. 2004; Jalaludin et al. 2007; Lepeule et al. 2010; Mannes et al. 2005; Pearce et al. 2010; Pesatori et al. 2008; Rich et al. 2009; Slama et al. 2009; van den Hooven et al. 2009).

PM concentration estimation. PM concentration estimates and estimation methods differed among the studies (Table 2). Some research groups relied on temporal variability in PM to estimate effects, where exposure was calculated by averaging all measurements over the entire study area for the pregnancy interval; for these studies, exposure estimates differed for pregnancies occurring at different times, but not by maternal residence, within the study area. Other studies estimated effects based on both temporal and spatial PM contrasts, where estimates were calculated for multiple geographic administrative units or at each maternal address; in these studies, exposures differed both by maternal address and by timing of the pregnancies within the study period. Most research groups (11 of 14; 79%) used routinely collected monitoring network data to estimate exposures (Table 2), although its use differs among studies [e.g., averages over geographic areas; nearest monitor measurement, or inverse distance-weighted (IDW) averages from multiple monitors, from residence].

Table 2: PM10 distribution, method of exposure<br />         estimation, area, and source of exposure variability, by study.

Table 2

PM10 distribution, method of exposure estimation, area, and source of exposure variability, by study.

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Two research groups used models to estimate PM10 exposure (Table 2), although modeling methods differed. The Generation R study (Rotterdam, the Netherlands) used dispersion modeling (combination of monitoring data with modeling techniques) (Wesseling et al. 2002), whereas the PIAMA study (Netherlands) used temporally adjusted land use regression (LUR) (Gehring et al. 2011) and estimated residential PM10 from modeled PM2.5 concentration (Cyrys et al. 2003). PAMPER used modeled estimates, as described above; the median modeled black smoke concentration in the PAMPER data set was 32.8 μg/m3 with an interquartile range of 17.1–104.9, reflecting, in part, the long time spanned. The Vancouver study used monitoring network data for PM10 but used both LUR models and monitoring network data (IDW) to estimate PM2.5 exposures (Brauer et al. 2008); results for both Vancouver PM2.5 estimates are shown below.

Socioeconomic status. Eleven of the 14 research groups used maternal education as the indicator of SES for model 1 (Table 1). However, the maternal education measure varied in form and meaning across studies. Three studies relied on contextual information based on neighborhood characteristics to define maternal SES for model 1 of the primary analysis (Table 1). Some research groups included additional individual level socioeconomic measures for model 2 and in secondary analyses [see Supplemental Material, Table 1 (doi:10.1289/ehp.1002725)]. For example, paternal occupation was used in the Lombardy study. The California study added area-level socioeconomic measures. Similarly, the Vancouver study added an additional area-level income variable. Some research groups included individual-level characteristics that may correlate with SES: maternal age, race, ethnicity, indigenous status, and country of birth.

Birth weight. Figure 1 shows the relative odds of term LBW per 10-μg/m3 increase in mean PM10 concentration during pregnancy, adjusted for SES (model 1) by location. Associations differed among study locations (p-value from test for heterogeneity < 0.001). Six studies indicated a statistically significant positive (adverse) association (Atlanta, California, Connecticut and Massachusetts, PAMPER, São Paulo, and Seoul), whereas the Sydney and Vancouver studies indicated an adverse, albeit not significant, association (Figure 1). Little or no association was reported by seven studies; no research group reported significant inverse (protective) associations.

Figure 1: ORs (95% CIs) for LBW among term births in association with a<br />         10‑μg/m3 increase in estimated average PM10, or black<br />         smoke (PAMPER), concentration during the entire pregnancy, adjusted for SES (model<br />         1), by study.

Figure 1

ORs (95% CIs) for LBW among term births in association with a 10‑μg/m3 increase in estimated average PM10, or black smoke (PAMPER), concentration during the entire pregnancy, adjusted for SES (model 1), by study.

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Figure 2 shows estimated ORs from model 2 [models fitted with additional covariates; see Supplemental Material, Table 1 (doi:10.1289/ehp.1002725)]. Additional covariates varied among studies and included maternal age and transformations of age, parity, antenatal visits, country of birth, sex, maternal smoking, maternal alcohol, maternal hypertension, maternal diabetes, season of conception, year of birth, marital status, race/ethnicity, indigenous status, gestational age, and contextual measures of SES. About half of model 2 ORs suggest slightly stronger associations between air pollution and term LBW compared with model 1 ORs, whereas other model 2 ORs were either very similar or attenuated compared with model 1 [for a direct comparison of estimates, see Supplemental Material, Table 2 (doi:10.1289/ehp.1002725). Associations differed among study locations (p-value from test for heterogeneity < 0.05).

Figure 2: ORs (95% CIs) for LBW among term births in association with a<br />         10‑μg/m3 increase in estimated average PM10, or black<br />         smoke (PAMPER), concentration during the entire pregnancy, adjusted for SES and<br />         study-specific variables (model 2), by study.

Figure 2

ORs (95% CIs) for LBW among term births in association with a 10‑μg/m3 increase in estimated average PM10, or black smoke (PAMPER), concentration during the entire pregnancy, adjusted for SES and study-specific variables (model 2), by study.

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Figure 3 shows changes in mean term birth weight associated with each 10-μg/m3 increase in PM10 for the 11 locations reporting continuous birth weight results. The mean estimated change ranged from a 42.2-g decrease (Generation R) to an increase of about 20 g (the Atlanta study), with most estimates (9 of 11) indicating a 2- to 20-g lower birth weight associated with each 10-μg/m3 increase in PM10 exposure. Of the 11 studies, six reported a statistically significant adverse effect of PM10, whereas two (the Atlanta and Lombardy studies) indicated a significant protective effect. These associations differed among study locations (p-value from test for heterogeneity < 0.001). After controlling for study-specific factors, model coefficients often, although not always, suggested larger decreases in birth weight with increases in PM10 [see Supplemental Material, Table 3 (doi:10.1289/ehp.1002725)]. In the Atlanta study, the estimate changed from an apparent mean increase of 20 g to a mean decrease of –28.8 g [95% confidence interval (CI), –49.6 to –8.1], whereas PIAMA’s estimate changed to an apparent increase [47.0 g (95% CI, –10.5 to 104.6)] after controlling for location-specific confounders.

Figure 3: Change in mean birth weight (95% CIs) among term births in<br />         association with a 10‑μg/m3 increase in estimated average<br />         PM10, or black smoke (PAMPER), concentration during the entire pregnancy,<br />         adjusted for SES, by study.

Figure 3

Change in mean birth weight (95% CIs) among term births in association with a 10‑μg/m3 increase in estimated average PM10, or black smoke (PAMPER), concentration during the entire pregnancy, adjusted for SES, by study.

Download larger image (TIF File)

Figure 4 shows estimated relative odds of LBW associated with each 10-μg/m3 increase in PM2.5 concentration, after controlling for SES, for a subset of studies. As for PM10, some studies indicated a significant increase in the relative odds of LBW, whereas others indicated no association. The Vancouver study reported different results using different PM2.5 estimates. p-Values from separate heterogeneity tests, each including one Vancouver estimate, were 0.06 (LUR) and 0.18 (IDW).

Figure 4: ORs (95% CIs) for LBW among term births in association with a<br />         10‑μg/m3 increase in estimated average PM2.5 concentration<br />         during the entire pregnancy, adjusted for SES, by study. Results for the Vancouver<br />         study are from two different PM2.5 estimation methods, LUR and IDW of<br />         monitor measurements (see "Methods").

Figure 4

ORs (95% CIs) for LBW among term births in association with a 10‑μg/m3 increase in estimated average PM2.5 concentration during the entire pregnancy, adjusted for SES, by study. Results for the Vancouver study are from two different PM2.5 estimation methods, LUR and IDW of monitor measurements (see “Methods”).

Download larger image (TIF File)


Despite the deliberately simple protocol and the heterogeneity in study designs and locations, we found some consistency across studies, particularly for the relationships between PM10 and mean birth weight and between PM2.5 and LBW. After controlling for SES, the reduction in mean birth weight associated with a PM10 increase of 10 μg/m3 was between 2 and 20 g for 9 of 11 locations. Although based on fewer studies than those for PM10, the initial tests of homogeneity for PM2.5 results were not statistically significant. More detailed meta-analysis of the initial results, considering alternative models, influential locations, and differences in location-specific covariates and exposures, may improve our understanding of these relationships and lead to improved summary estimates.

Based on a discussion of initial feasibility study results at the 2009 workshop in Dublin, Ireland (see Appendix), participants concluded that the method used to estimate PM10 exposures may be the most critical design difference among the studies. Some prior studies from California (Basu et al. 2004; Wilhelm and Ritz 2005), Vancouver (Brauer et al. 2008), Sydney (Mannes et al. 2005), and Atlanta (Darrow et al. 2009a) have examined the consequences of different methods for calculating pollution metrics in the same study but from different perspectives. For example, as in the results presented in Figure 4, Brauer et al. (2008) compared PM2.5 estimates from LUR and monitor data (IDW) and concluded that their moderate correlation could be attributable to different aspects of variability being captured by each method. Basu et al. (2004) found stronger associations for exposures estimated over larger geographic areas than over smaller geographic areas but did not speculate on the reasons for the discrepancy; however, Basu et al. (2004) cautioned that studies using different methods for exposure assessment may not be comparable.

Importantly, there is large variation in PM10 levels and concentration ranges among study locations. In the Vancouver study, for example, the 10-μg/m3 increase used to derive ORs is nearly an order of magnitude greater than the interquartile range (11.7–13.1; Table 2) of exposures. Similarly, in the Atlanta study, the 10-μg/m3 reporting unit represents nearly the entire range of PM10 concentrations (18.6–29.6 μg/m3).The analytical methods used in the common framework assume no threshold level below which PM is not associated with health. Although evidence supports the hypothesis that no threshold exists for PM relationships and overall population mortality (Daniels et al. 2000), threshold assumptions have not been fully explored for adverse reproductive outcomes, including birth weight. We did not directly examine nonlinear relationships in this feasibility study, but they may contribute to heterogeneity among studies; a more fully coordinated analysis should improve our ability to assess nonlinear relationships.

Covariates likely to affect the relationship between PM10 and LBW differ among study locations for many reasons (Strickland et al. 2009). For studies that estimate effects based on spatial contrasts, controlling for SES can be important because it may be spatially correlated with exposure concentrations (O’Neill et al. 2003). However, SES measures and their relationships with both birth outcomes and air pollution are not consistent. For example, although mothers with lower SES generally tend to have poorer birth outcomes, the strength of the relationship differs depending on which birth outcome (birth weight, preterm birth) and which measures of SES (maternal education, occupation) are used (Parker et al. 1994; Pickett et al. 2002). Although in some places mothers with higher SES live in less-polluted areas (Woodruff et al. 2003), in others the opposite relationship holds (Slama et al. 2007). Because participating studies rely on exposure estimates with differing spatial and temporal components, critical confounders may differ among studies (Strickland et al. 2009). Changes between results for the models using SES only and those using SES plus covariates varied among studies, suggesting that other statistical approaches, possibly hierarchical models, that allow for different types of confounding factors could be informative for understanding apparent variations among locations.

Finally, other methods of analysis could be used. Although logistic regression is commonly applied, alternative approaches have considered spatial correlations (Jerrett et al. 2005), time-varying exposures (Suh et al. 2009), generalized additive models (Ballester et al. 2010), and hierarchical structures (Yi et al. 2010). Bell et al. (2007) proposed a method for handling correlated exposures across trimesters. Because both model-based and spatially averaged exposure estimates are calculated with error, considering their precision would provide more accurate confidence intervals (Woodruff et al. 2009).

The ICAPPO feasibility project successfully coordinated analyses of the association between ambient PM concentrations and term LBW, across multiple locations, data sets, and research teams worldwide. These initial results and the participation of multiple research groups, even without external funding, support the continuation of this effort to increase our understanding of the human reproductive consequences of adverse air quality.


We thank Jason Harless for coordinating many aspects of the feasibility study and all of the participants at the 2009 Dublin, Ireland, ICAPPO workshop who contributed their insights and ideas: I. Aguilera, F. Ballester, K. Belanger, M.-H.Chang, G. Collman, M. Dostal, K. Gray, C. Iñiguez, B.-M. Kim, K. Polanska, and J. Rankin.

We thank the principal investigators and scientific teams of the participating centers. For the PIAMA study: B. Brunekreef (Utrecht University and University Medical Center Utrecht, the Netherlands); H.A. Smit [National Institute for Public Health and the Environment (RIVM) and University Medical Center Utrecht, the Netherlands]; A.H. Wijga (RIVM, the Netherlands); J.C. de Jongste (Erasmus University Medical Center/Sophia Children’s Hospital Rotterdam, the Netherlands); J. Gerritsen, D.S. Postma, M. Kerkhof, and G.H. Koppelman (Medical Center Groningen, the Netherlands); and R.C. Aalberse (Sanquin Research, Amsterdam, the Netherlands). The PIAMA study is supported by the Netherlands Organization for Health Research and Development; the Netherlands Organization for Scientific Research; the Netherlands Asthma Fund; the Netherlands Ministry of Spatial Planning, Housing, and the Environment; and the Netherlands Ministry of Health, Welfare, and Sport. For the PAMPER study: L. Parker (Dalhousie University, Halifax, Nova Scotia, Canada) and T. Pless-Mulloli (Newcastle University, Newcastle upon Tyne, United Kingdom). The PAMPER study was supported by the Wellcome Trust (grant No 072465/Z/03/Z). For the Eden study: M.-A. Charles and her group (INSERM 1018 and INSERM–INED joint research team).

For the Vancouver analysis, the linked research database was provided by Population Data BC. Medical services and hospitalization data were provided by the Ministry of Health, Government of British Columbia; Vital Statistics data, by the British Columbia Vital Statistics Agency; and perinatal data, by the British Columbia Reproductive Care Program.


  1. Australian Bureau of Statistics 2001. Socio-economic Indexes for Areas, Australia 2001. ABS Catalogue no. 2039.0. Canberra:Australian Bureau of Statistics.
  2. Baccarelli A, Zanobetti A, Martinelli I, Grillo P, Hou L, Lanzani G, et al. 2007. Air pollution, smoking, and plasma homocysteine. Environ Health Perspect 115:176–181.
  3. Ballester F, Estarlich M, Iñiguez C, Llop S, Ramón R, Esplugues A, et al. 2010. Air pollution exposure during pregnancy and reduced birth size: a prospective birth cohort study in Valencia, Spain. Environ Health 9:6.doi:10.1186/1476-069X-9-6
  4. Basu R, Woodruff TJ, Parker JD, Saulnier L, Schoendorf KC. 2004. Comparing exposure metrics in the relationship between PM2.5 and birth weight in California. J Expo Anal Environ Epidemiol 14:391–396.
  5. Bell ML, Ebisu K, Belanger K. 2007. Ambient air pollution and low birth weight in Connecticut and Massachusetts. Environ Health Perspect 115:1118–1125.
  6. Bell ML, Ebisu K, Belanger K. 2008. The relationship between air pollution and low birth weight: effects by mother’s age, infant sex, co-pollutants, and pre-term births. Environ Res Lett 3:044003.doi: 10.1088/1748-9326/3/4/044003
  7. Brauer M, Lencar C, Tamburic L, Koehoorn M, Demers P, Karr C.. 2008. A cohort study of traffic-related air pollution impacts on birth outcomes. Environ Health Perspect 116:680–686.
  8. Cyrys J, Heinrich J, Hoek G, Meliefste K, Lewne M, Gehring U, et al. 2003. Comparison between different particle indicators: elemental carbon (EC), PM2.5 mass and absorbance. J Expo Anal Environ Epidemiol 13:134–143.
  9. Daniels MJ, Dominici F, Samet JM, Zeger SL. 2000. Estimating particulate matter-mortality dose-response curves and threshold levels: an analysis of daily time series for the 20 largest US cities. Am J Epidemiol 152:397–406.
  10. Darrow LA, Klein M, Flanders WD, Waller LA, Correa A, Marcus M, et al. 2009. . Ambient air pollution and preterm birth: a time-series analysis. Epidemiology 20:689–698.
  11. Darrow LA, Strickland MJ, Klein M, Waller LA, Flanders WD, Correa A, et al. 2009. . Seasonality of birth and implications for temporal studies of preterm birth. Epidemiology 20:699–706.
  12. Fanshawe TR, Diggle PJ, Rushton S, Sanderson R, Lurz PWW, Glinianaia SV, et al. 2008. Modelling spatio-temporal variation in exposure to particulate matter: a two-stage approach. Environmetrics 19:549–566.
  13. Gehring U, Wijga AH, Fischer P, de Jongste JC, Kerkhof M, Koppelman GH, et al. 2011. Traffic-related air pollution, preterm birth and term birth weight in the PIAMA birth cohort study. Environ Res 111(1):125–135.
  14. Glinianaia SV, Rankin J, Bell R, Pless-Mulloli T, Howel D. 2004. Particulate air pollution and fetal health: a systematic review of the epidemiologic evidence. Epidemiology 15:36–45.
  15. Glinianaia SV, Rankin J, Pless-Mulloli T, Pearce MS, Charlton M, Parker L. 2008. Temporal changes in key maternal and fetal factors affecting birth outcomes: a 32-year population-based study in an industrial city. BMC Pregnancy Childbirth 8:39.doi: 10.1186/1471-2393-8-39
  16. Gouveia N, Bremner SA, Novaes HM. 2004. Association between ambient air pollution and birth weight in São Paulo, Brazil. J Epidemiol Community Health 58:11–17.
  17. Ha EH, Lee BE, Park HS, Kim YS, Kim H, Kim YJ, et al. 2004. Prenatal exposure to PM10 and preterm birth between 1998 and 2000 in Seoul, Korea. J Prev Med Public Health 37:300–305.
  18. Ivy D, Mulholland J, Russell A.. 2008. Development of ambient air quality population-weighted metrics for use in time-series health studies. J Air Waste Manag Assoc 58:711–720.
  19. Jalaludin B, Mannes T, Morgan G, Lincoln D, Sheppeard V, Corbett S.. 2007. Impact of ambient air pollution on gestational age is modified by season in Sydney, Australia. Environ Health 6:16.doi:10.1186/1476-069X-6-16
  20. Jerrett M, Burnett RT, Ma R, Pope CA III, Krewski D, Newbold KB, et al. 2005. Spatial analysis of air pollution and mortality in Los Angeles. Epidemiology 16:727–736.
  21. Kaufman JS, Alonso FT, Pino P. 2008. Multi-level modeling of social factors and preterm delivery in Santiago de Chile. BMC Pregnancy Childbirth 8:46..
  22. Lepeule J, Caini F, Bottagisi S, Galineau J, Hulin A, Marquis N, et al. 2010. Maternal exposure to nitrogen dioxide during pregnancy and offspring birth weight: comparison of two exposure models. Environ Health Perspect 118:1483–1489.
  23. Mannes T, Jalaludin B, Morgan G, Lincoln D, Sheppeard V, Corbett S.. 2005. Impact of ambient air pollution on birth weight in Sydney, Australia. Occup Environ Med 62:524–530.
  24. Morello-Frosch R, Jesdale BM, Sadd JL, Pastor M. 2010. Ambient air pollution exposure and full-term birth weight in California. Environ Health 9:44.doi:10.1186/1476-069X-9-44
  25. Muir D, Laxen DP. 1995. Black smoke as a surrogate for PM10 in health studies. Atmos Environ 29:959–962.
  26. O’Neill MS, Jerrett M, Kawachi I, Levy JI, Cohen AJ, Gouveia N, et al. 2003. Health, wealth, and air pollution: advancing theory and methods. Environ Health Perspect 111:1861–1870.
  27. Parker JD, Schoendorf KC, Kiely JL. 1994. Associations between measures of socioeconomic status and low birth weight, small for gestational age, and premature delivery in the United States. Ann Epidemiol 4:271–278.
  28. Pearce MS, Glinianaia SV, Rankin J, Rushton S, Charlton M, Parker L, et al. 2010. No association between ambient particulate matter exposure during pregnancy and stillbirth risk in the north of England, 1962–1992. Environ Res 110:118–122.
  29. Pesatori AC, Bonzini M, Carugno M, Giovannini N, Signorelli V, Baccarelli A, et al. 2008. Ambient air pollution affects birth and placental weight. A study from Lombardy (Italy) region. Epidemiology 19: suppl178–179.
  30. Pickett KE, Ahern JE, Selvin S, Abrams B. 2002. Neighborhood socioeconomic status, maternal race and preterm delivery: a case-control study. Ann Epidemiol 12:410–418.
  31. Rich DQ, Demissie K, Lu SE, Kamat L, Wartenberg D, Rhoads GG. 2009. Ambient air pollutant concentrations during pregnancy and the risk of fetal growth restriction. J Epidemiol Community Health 63:488–496.
  32. Ritz B, Wilhelm M.. 2008. Ambient air pollution and adverse birth outcomes: methodologic issues in an emerging field. Basic Clin Pharmacol Toxicol 102:182–190.
  33. Slama R, Darrow L, Parker J, Woodruff TJ, Strickland M, Nieuwenhuijsen M, et al. 2008. Meeting report: atmospheric pollution and human reproduction. Environ Health Perspect 116:791–798.
  34. Slama R, Morgenstern V, Cyrys J, Zutavern A, Herbarth O, Wichmann HE, et al. 2007. Traffic-related atmospheric pollutants levels during pregnancy and offspring’s term birth weight: a study relying on land-use-regression exposure models. Environ Health Perspect 115:1283–1292.
  35. Slama R, Thiebaugeorges O, Goua V, Aussel L, Sacco P, Bohet A, et al. 2009. Maternal personal exposure to airborne benzene and intrauterine growth. Environ Health Perspect 117:1313–1321.
  36. Šrám RJ, Binková B, Dejmek J, Bobak M. 2005. Ambient air pollution and pregnancy outcomes: a review of the literature. Environ Health Perspect 113:375–382.
  37. Sterne JAC, Bradburn MJ, Egger M. 2001. Meta-analysis in Stata. In: Systematic Reviews in Health Care: Meta-Analysis in Context, 2nd ed. (Egger M, Davey Smith G, Altman DA, eds). London:BMJ Publishing. pp. 347–369.
  38. Strickland MJ, Klein M, Darrow LA, Flanders WD, Correa A, Marcus M, et al. 2009. The issue of confounding in epidemiological studies of ambient air pollution and pregnancy outcomes. J Epidemiol Community Health 63:500–504.
  39. Suh YJ, Kim H, Seo JH, Park H, Kim YJ, Hong YC, et al. 2009. Different effects of PM10 exposure on preterm birth by gestational period estimated from time-dependent survival analyses. Int Arch Occup Environ Health 82:613–621.
  40. Townsend P, Phillimore P, Beattie A. 1988. Health and Deprivation: Inequality and the North. London:Routledge.
  41. van den Hooven EH, Jaddoe VW, de Kluizenaar Y, Hofman A, Mackenbach JP, Steegers EA, et al. 2009. Residential traffic exposure and pregnancy-related outcomes: a prospective birth cohort study. Environ Health 8:59.doi:10.1186/1476-069X-8-59
  42. Wesseling J, den Boeft J, Boersen GAC, Hollander K, van den Hout KD, Keuken MP, et al. Development and validation of the new TNO model for the dispersion of traffic emissions. In: 8th International Conference on Harmonisation within Atmospheric Dispersion Modelling for Regulatory Purposes.; Sofia, Bulgaria:Demetra Ltd.. 2002. pp. 456–460.
  43. Wilhelm M, Ritz B.. 2005. Local variations in CO and particulate air pollution and adverse birth outcomes in Los Angeles County, California, USA. Environ Health Perspect 113:1212–1221.
  44. Woodruff TJ, Parker JD, Adams K, Bell ML, Gehring U, Glinianaia S, et al. 2010. International Collaboration on Air Pollution and Pregnancy Outcomes (ICAPPO). Int J Environ Res Public Health 7:2638–2652.
  45. Woodruff TJ, Parker JD, Darrow LA, Slama R, Bell ML, Choi H, et al. 2009. Methodological issues in studies of air pollution and reproductive health. Environ Res 109:311–320.
  46. Woodruff TJ, Parker JD, Kyle AD, Schoendorf KC. 2003. Disparities in exposure to air pollution during pregnancy. Environ Health Perspect 111:942–946.
  47. Yi O, Kim H, Ha E.. 2010. Does area level socioeconomic status modify the effects of PM10 on preterm delivery? Environ Res 110:55–61.

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